EP4213162A1 - Procédé d'élimination de radionucléides de déchets radioactifs aqueux - Google Patents

Procédé d'élimination de radionucléides de déchets radioactifs aqueux Download PDF

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Publication number
EP4213162A1
EP4213162A1 EP22153522.2A EP22153522A EP4213162A1 EP 4213162 A1 EP4213162 A1 EP 4213162A1 EP 22153522 A EP22153522 A EP 22153522A EP 4213162 A1 EP4213162 A1 EP 4213162A1
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EP
European Patent Office
Prior art keywords
radioactive waste
waste solution
precipitate
aqueous
zirconium
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EP22153522.2A
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German (de)
English (en)
Inventor
Sumit PAHAN
Arvind ANANTHANARAYANAN
Raman Kumar Mishra
Dayamoy Banerjee
Tessy VINCENT
Sugilal Gopalakrishnan
Chetan Parkash Kaushik
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Secretary Department Of Atomic Energy Government Of India
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Secretary Department Of Atomic Energy Government Of India
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Publication of EP4213162A1 publication Critical patent/EP4213162A1/fr
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    • G—PHYSICS
    • G21—NUCLEAR PHYSICS; NUCLEAR ENGINEERING
    • G21F—PROTECTION AGAINST X-RADIATION, GAMMA RADIATION, CORPUSCULAR RADIATION OR PARTICLE BOMBARDMENT; TREATING RADIOACTIVELY CONTAMINATED MATERIAL; DECONTAMINATION ARRANGEMENTS THEREFOR
    • G21F9/00—Treating radioactively contaminated material; Decontamination arrangements therefor
    • G21F9/04—Treating liquids
    • G21F9/06—Processing
    • G21F9/10—Processing by flocculation
    • G—PHYSICS
    • G21—NUCLEAR PHYSICS; NUCLEAR ENGINEERING
    • G21F—PROTECTION AGAINST X-RADIATION, GAMMA RADIATION, CORPUSCULAR RADIATION OR PARTICLE BOMBARDMENT; TREATING RADIOACTIVELY CONTAMINATED MATERIAL; DECONTAMINATION ARRANGEMENTS THEREFOR
    • G21F9/00—Treating radioactively contaminated material; Decontamination arrangements therefor
    • G21F9/04—Treating liquids
    • G21F9/06—Processing
    • G21F9/12—Processing by absorption; by adsorption; by ion-exchange
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/52—Treatment of water, waste water, or sewage by flocculation or precipitation of suspended impurities
    • C02F1/5236—Treatment of water, waste water, or sewage by flocculation or precipitation of suspended impurities using inorganic agents
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/58—Treatment of water, waste water, or sewage by removing specified dissolved compounds
    • C02F1/62—Heavy metal compounds
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/66—Treatment of water, waste water, or sewage by neutralisation; pH adjustment
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F1/00—Treatment of water, waste water, or sewage
    • C02F1/68—Treatment of water, waste water, or sewage by addition of specified substances, e.g. trace elements, for ameliorating potable water
    • G—PHYSICS
    • G21—NUCLEAR PHYSICS; NUCLEAR ENGINEERING
    • G21F—PROTECTION AGAINST X-RADIATION, GAMMA RADIATION, CORPUSCULAR RADIATION OR PARTICLE BOMBARDMENT; TREATING RADIOACTIVELY CONTAMINATED MATERIAL; DECONTAMINATION ARRANGEMENTS THEREFOR
    • G21F9/00—Treating radioactively contaminated material; Decontamination arrangements therefor
    • G21F9/04—Treating liquids
    • G21F9/06—Processing
    • G21F9/12—Processing by absorption; by adsorption; by ion-exchange
    • G21F9/125—Processing by absorption; by adsorption; by ion-exchange by solvent extraction
    • C—CHEMISTRY; METALLURGY
    • C02—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F—TREATMENT OF WATER, WASTE WATER, SEWAGE, OR SLUDGE
    • C02F2101/00—Nature of the contaminant
    • C02F2101/006—Radioactive compounds

Definitions

  • the present invention relates to the field of radioactive waste (IPC class G21C 19/00), specifically to a method for the separation of radionuclides from an aqueous radioactive waste solution management (IPC class G21C 19/46).
  • the present invention also relates to a corresponding use.
  • Radionuclides are significant dose contributors in radioactive waste, especially in intermediate level radioactive Waste (ILW) and low level radioactive waste (LLW).
  • ILW intermediate level radioactive Waste
  • LLW low level radioactive waste
  • a present strategy for the management of these species/elements is a delay and decay approach with the intermediate level waste held in tanks for the period of around 30 years prior to discharge. However, this adds greatly to the cost of intermediate level radioactive waste and low level radioactive waste management at the back end of the fuel cycle of a nuclear power plant.
  • EP 2 224 354 7 A1 discloses a sorbent for antimony anions, consisting essentially of particles or granules of zirconium oxide having a distribution coefficient for antimony anions of at least 10,000 ml/g.
  • the disadvantage of this sorbent is that it is not water soluble and that only antimony are targeted while ruthenium ions are not addressed in the disclosure.
  • EP 3 396 677 A1 also discloses a solid adsorbent capable of adsorbing radioactive antimony, radioactive iodine and radioactive ruthenium, the adsorbent comprising cerium (IV) hydroxide, wherein the cerium (IV) hydroxide has the following properties: (1) a granular form having a particle size of 250 ⁇ m or more and 1200 ⁇ m or less, (2) in a thermogravimetric analysis, a weight reduction ratio is 4.0% or more and 10.0% or less when the temperature is increased from 200 °C to 600 °C, and (3) in an infrared absorption spectrum analysis, absorption peaks are observed in ranges of 3270 cm -1 or more and 3330 cm -1 or less, 1590 cm -1 or more and 1650 cm -1 or less, and 1410 cm -1 or more and 1480 cm -1 or less.
  • This method has also the disadvantage, that a solid adsorbent media has to be provided, through which a nuclear wastes passes through.
  • the objective behind the present invention is thus the development of a process for the removal of radionuclides from an aqueous radioactive waste solution to significantly reduce the volume of radioactive waste to lower the environmental and economic footprint associated with aqueous radioactive waste management.
  • a method for the separation of radionuclides from an aqueous radioactive waste solution comprising:
  • the pH change results in the precipitation of various iron hydroxides and iron oxyhydroxides, which can adsorb radionuclides. It was surprisingly found that the use of zirconium salts increases the efficiency of the adsorption process.
  • the method further comprises flocculating the precipitate P, after the changing of the pH. Flocculating can help to increase the particle size of the precipitated species after changing of the pH, which can be beneficial for an efficient separation of the precipitate P from the radioactive waste solution.
  • Aspect three according to the first or second aspect of the present invention discloses a method further comprising, processing the solution obtained after separating the precipitate P to remove further species, preferably cesium and strontium species, prior to discharge. It can be necessary to further treat the radioactive waste solution obtained after separating the precipitate P to lower the environmental and health hazards prior to discharge. To this regard, the removal of cytotoxic cesium and strontium can be mandatory prior to discharging to the treated radioactive waste solution.
  • a method is disclosed, wherein the at least one zirconium salt is added to the received aqueous radioactive waste solution prior to changing the pH of the radioactive waste solution to obtain the precipitate P.
  • the at least one zirconium salt is added to the received aqueous radioactive waste solution after changing the pH of the radioactive waste solution to obtain the precipitate P.
  • the zirconium salt added to the aqueous radioactive waste solution is selected from zirconium salts with zirconium ions having an oxidation level of +4, preferably from the group comprising zirconium oxychloride, zirconium nitrate or a zirconium oxynitrate or any mixture thereof. It was found that these zirconium slats allow for high decontamination factors.
  • the decontamination factor is calculated by dividing the specific activity of the radionuclides in Becquerel/milliliter in the provided aqueous radioactive waste by the activity of radionuclides in Becquerel/milliliter of the obtained aqueous solution after separating the precipitate P from the radioactive waste solution.
  • zirconium slats being particular efficient in decreasing the decontamination factor, also other water soluble zirconium salts can be used.
  • the at least one zirconium salt is added in its solid form and/or as an aqueous solution comprising the at least one zirconium salt.
  • a solution of the at least one zirconium salt can be added to the radioactive waste solution.
  • the addition of the at least one zirconium salt is added in its solid form also ensures the efficient removal of radionuclides after the pH change.
  • the zirconium concentration of the solution obtained after adding at least one zirconium salt to the aqueous radioactive waste solution is in the range of 0.5 to 2.5 mg/l zirconium, preferably 1.0 to 2.25 mg/l zirconium, most preferably 1.5 to 2.0 mg/l. It was found, that a certain zirconium concentration needs to be exceeded to achieve high decontamination factors for the radioactive waste solution
  • the pH of the of the radioactive waste solution is changed to a pH range of 6 to 8, preferably to a pH of 6.5 to 7.5.
  • the method is less efficient at an alkaline pH due to blocking of surface-active sites by hydroxide ions (OH - ) from the solution.
  • the process works most efficiently at near neutral pH (pH 6 to 8).
  • the aqueous radioactive waste contains significant concentrations of iron based corrosion products arising from the degradation of piping and other plant components. When the pH is changed towards the neutral region, most of these iron based corrosion products precipitate as iron hydroxides and oxyhydroxides.
  • the aqueous radioactive waste solution is an acidic or alkaline intermediate or low level radioactive waste solution, preferably an acidic intermediate and/or low level radioactive waste solution.
  • the process is most suitable for acidic intermediate or low level radioactive waste. It works also for alkaline intermediate or low level radioactive waste but with reduced efficiency. The reduced efficiency at an alkaline pH is most likely caused by blocking of surface-active sites by hydroxide ions (OH - ) from the solution.
  • the difference between low level and intermediate level radioactive waste is essentially only the activity of the waste and not the composition of the solution itself.
  • the difference between acidic and alkaline radioactive waste is essentially only the pH of the radioactive waste solution.
  • the activity of intermediate level radioactive waste is considered to range from around 3.7 ⁇ 10 ⁇ 4 Bq/ml to around 3.7 ⁇ 10 ⁇ 7 Bq/ml and low level radioactive waste therefore has an activity of less than around 3.7 ⁇ 10 ⁇ 4 Bq/ml.
  • the pH of the of the radioactive waste solution is changed by adding at least one additive in the form of a base to the received acidic aqueous low or intermediate level radioactive waste solution.
  • the pH of the radioactive waste solution is changed by adding at least one additive in the form of an acid to the received alkaline low or intermediate level radioactive waste solution.
  • the at least one base is a water soluble salt and/or an aqueous solution of a water soluble salt
  • the water soluble salt is preferably an alkali metal hydroxide, more preferably sodium hydroxide, potassium hydroxide, lithium hydroxide, rubidium hydroxide, wherein sodium hydroxide is preferred or the at least one acid is hydrochloric acid (HCl), nitric acid (HNO 3 ) or sulfuric acid (H 2 SO 4 ), wherein 1 M nitric acid is preferred.
  • an aqueous solution of the at least one base can be added to the radioactive waste solution.
  • the addition of the at least on base in its solid form also ensures the efficient removal of radionuclides after the pH change. Strong bases like alkali metal hydroxides are preferred to limit the amount of mass added to the radioactive waste solution.
  • Radionuclides comprise ruthenium isotopes, preferably with a mass number of 106 and antimony isotopes, preferably with a mass number of 125. Both elements are significant dose contributors in radioactive waste, especially acidic intermediate or low level radioactive waste.
  • Aspect fourteen of the present invention discloses a method, wherein the precipitate P comprises or consists of ruthenium and/or antimony, preferably and wherein ruthenium and/or antimony are precipitated simultaneously.
  • the method according to the invention it is possible to simultaneously separate both ruthenium and antimony radionuclides. Simultaneous precipitation of both species allows for a single step precipitation which results in a cost effective method for the treatment of radioactive waste.
  • the separation of the precipitate P from the radioactive waste solution comprises the filtration or centrifugation of the solution obtained after changing the pH of the radioactive waste solution to obtain a precipitate P or flocculating the precipitate P, after the changing of the pH.
  • the relatively small volume of radionuclides bearing precipitates after their separation can be easily handled final storage in e.g. a solid cement block or similar matrices for final storage of the radioactive waste, which greatly reduces space requirements and cost for the management of radioactive waste. Since the precipitation and filtration occurs directly in the liquid, further steps necessary to fabricate/synthesize a supported sorbent structure is prevented. This aids in simplicity for scale-up, while maintaining high surface activity inherent in the solution state.
  • the activity in Becquerel/milliliter caused by ruthenium 106 and antimony 125 in the supernatant obtained after process step e) is at least 20 times, preferably 100, more preferably at least 300 times, even more preferably 500 times lower than the activity of the received aqueous radioactive waste solution, and wherein the activity in Becquerel/milliliter caused by ruthenium 106 and antimony 125 in the supernatant obtained after separating the precipitate P from the acidic radioactive waste solution is at least 100 times, preferably 300, more preferably at least 500 times lower than the activity of the received aqueous radioactive waste solution, and wherein the activity in Becquerel/milliliter caused by ruthenium 106 and antimony 125 in the supernatant obtained after separating the precipitate P from the alkaline radioactive waste solution is at least 20 times, preferably 30 times lower than the activity of the received aqueous radioactive waste
  • the activity in Becquerel/milliliter caused by ruthenium 106 and antimony 125 in the supernatant obtained after process step e) is at least 20 times, preferably 100, more preferably at least 300 times, even more preferably 500 times lower than the activity of the received aqueous radioactive waste solution, or wherein the activity in Becquerel/milliliter caused by ruthenium 106 and antimony 125 in the supernatant obtained after separating the precipitate P from the acidic radioactive waste solution is at least 100 times, preferably 300, more preferably at least 500 times lower than the activity of the received aqueous radioactive waste solution, or wherein the activity in Becquerel/milliliter caused by ruthenium 106 and antimony 125 in the supernatant obtained after separating the precipitate P from the alkaline radioactive waste solution is at least 20 times, preferably 30 times lower than the activity of the received aqueous radio
  • aspects nineteen of the present invention discloses the use of zirconium salts, preferably zirconium oxychloride, zirconium nitrate or a zirconium oxynitrate or any mixture thereof, for the treatment of aqueous radioactive waste solution, preferably acidic or alkaline intermediate or low level radioactive waste solution, preferably an acidic intermediate and/or low level radioactive waste solution.
  • aqueous radioactive waste solution preferably acidic or alkaline intermediate or low level radioactive waste solution, preferably an acidic intermediate and/or low level radioactive waste solution.
  • the method according to the invention is directed to the separation of radionuclides form aqueous radioactive waste by adding soluble salts of zirconium to the aqueous radioactive waste and conducting a single pH-changing step.
  • the radionuclides bearing precipitates can be separated to obtain a clean, radionuclides lean solution.
  • This radionuclides lean solution can then be subjected to further treatments as necessary prior to discharge.
  • the relatively small volume of precipitates can be isolated, which greatly reduces space requirements and costs, which allows significant reductions in the ecological and economic footprint of radioactive waste management.
  • a method for the separation of radionuclides from an aqueous radioactive waste solution comprising: a) receiving of an aqueous radioactive waste solution, b) adding at least one zirconium salt to the aqueous radioactive waste solution, c) changing the pH of the radioactive waste solution to obtain a precipitate P, and d) separating the precipitate P from the radioactive waste solution.
  • FIG. 1 shows a flow chart of the method according an embodiment of the present invention.
  • aqueous radioactive waste solution is received.
  • the at least one zirconium salt is added to the aqueous radioactive waste solution.
  • the pH of the radioactive waste solution is changed to obtain a precipitate P.
  • the precipitate P is separated from the radioactive waste solution. It can also be possible to change the pH of the radioactive waste solution prior to adding the at least one zirconium salt, meaning that step c) is conducted before step b).
  • the operations of the method can be especially effective in an in-situ process for the separation of the radionuclides ruthenium 106 and antimony 125 from acidic intermediate level radioactive waste and low level radioactive waste.
  • Ruthenium 106 and antimony 125 constitute a significant hazard in intermediate level radioactive waste and low level radioactive waste management, as they are radiotoxic and cytotoxic.
  • a pH change results in the precipitation of various iron hydroxides and iron oxyhydroxides, which can adsorb radionuclides, in particular ones like ruthenium and antimony.
  • the inventors have recognized that the use of zirconium salts increases the efficiency of the adsorption process.
  • FIG. 2 illustrates a preferred embodiment of the present invention for the simultaneous removal of ruthenium and antimony from acidic intermediate level radioactive waste (ILW), comprising the steps:
  • a ruthenium 106 and antimony 125 bearing phase of much smaller volume than the original provided acidic aqueous intermediate level radioactive waste can be stored for further processing.
  • the decontamination factor (DF) for Ruthenium 106 and Antimony 125 significantly exceeds 300, so that the intermediate level radioactive waste can be discharged after cesium and strontium removal.
  • Table 1 A detailed waste composition which is treated with the method according to the invention.
  • Typical characteristics of acidic raffinate post PUREX, actinide and fission product removal HNO 3 molarity (M) 3.7 Gross ⁇ radiation (Bq/ml) 21 Gross Beta radiation (Bq/ml) 4.4 ⁇ 10 5 137 Cs (Bq/ml) 4.1 ⁇ 10 3 90 Sr & 90 Y (Bq/ml) ⁇ 4.1 ⁇ 10 3 134 Cs (Bq/ml) ⁇ 4.1 ⁇ 10 3 125 Sb (Bq/ml) 2.2 ⁇ 10 5 - 3.0 ⁇ 10 5 106 Ru (Bq/ml) 7.4 ⁇ 10 4 - 1.1 ⁇ 10 5
  • PUREX means that plutonium-uranium recovery by extraction was already aqueous radioactive waste, as well as actinide and fission product removal.
  • Decontamination factor DF Activity of the received radioactive waste solution
  • the detection was performed by gamma spectroscopy using a calibrated multi-channel analyzer (MCA) to detect the 428 keV gamma emission of antimony 125 and 511 keV gamma emission of ruthenium 106.
  • MCA multi-channel analyzer
  • 0.5 ml of the solution to be analyzed were taken in a gamma vial and placed in the analyzer for measurement.
  • the higher activity wastes were measured for around 10 minutes, while the low activity solutions, e.g. the solution after precipitation and separation of the ruthenium and antimony species, required hour of measurement to accumulate enough data. Each measurement was repeated at least three times to ensure accuracy.
  • the limit of detection with the applied gamma spectroscopy is around 19 Bq/ml.
  • Example 1 Effect of pH on ruthenium 106 and antimony 125 removal by in-situ precipitation of zirconium (IV) hydroxide (Zr(OH) 4 ).
  • the first batch of studies were carried out on a 50 ml scale using cesium lean intermediate level radioactive waste to ascertain the effect of pH on ruthenium and antimony removal.
  • Table 1 a constant zirconium dosing of 1.0 mg/l zirconyl dichloride (ZrOCl 2 ) was maintained. Starting pH was varied between 4 to 12.
  • Ruthenium 106 activity in the feed was 9.6 ⁇ 10 4 Bq/ml, while antimony125 activity was 2.3 ⁇ 10 5 Bq/ml.
  • Table 2 summarizes the effect of pH on the decontamination factor.
  • Table 2 Effect of the pH on the Ruthenium 106 and Antimony 125 decontamination factor. pH Decontamination factor of antimony 125 Supernatant activity of ruthenium 106 4 415 342 6 1000 below limit of detection 8 810 1368 10 270 162 12 220 13
  • Table 2 shows that the Decontamination Factor (DF) obtained are highest for both antimony and ruthenium between pH 6 to 8, indicating that the process works most optimally at circumneutral pH.
  • Example 2 Effect of the zirconium concentration on ruthenium and antimony removal by in-situ precipitation of zirconium hydroxide (Zr(OH) 4 ).
  • Zr(OH) 4 zirconium hydroxide
  • the concentration of zirconium in the solution obtained using zirconyl dichloride (ZrOCl 2 ) was varied at a constant pH of 6 of the solution and the effect on ruthenium and antimony removal was observed.
  • Ruthenium 106 activity in the feed was 9.6 Bq/ml, while antimony 125 activity was 2.3 ⁇ 10 5 Bq/ml.
  • Table 3 Effect of the zirconium concentration on the ruthenium 106 and antimony 125 decontamination factor according to example 2.
  • zirconium concentrations of 2.0 mg/l or greater allows most efficient removal of ruthenium 106 and antimony 125.
  • Example 3 Effect of zirconium source on ruthenium 106 and antimony125removal by in-situ precipitation of zirconium (IV) hydroxide (Zr(OH) 4 ).
  • zirconium (IV) hydroxide (Zr(OH) 4 ) The effect of various zirconium sources to achieve a zirconium concentration of 1.0 mg/l in the acidic intermediate level radioactive waste at pH 6 was investigated. Ruthenium106 activity in the feed was 2.1 Bq/ml, while antimony 125 activity was 9.5 Bq/ml. The results of these studies are collected in Table 4.
  • Table 4 Effect of zirconium source on ruthenium 106 and antimony 125 removal according to example 3.
  • Example 4 Decontamination factors achieved for intermediate alkaline radioactive waste with a pH of 12.
  • concentration of zirconium in the solution obtained using zirconyl dichloride (ZrOCl 2 ) was adjusted to 1.0 mg/l, followed by the addition of 1 M nitric acid to reduce the pH of the radioactive waste solution to pH 6 to 7.
  • Ruthenium 106 activity in the feed was 9.6 Bq/ml, while antimony 125 activity was 2.5 ⁇ 10 5 Bq/ml.
  • Table 5 Effect on the activity of intermediate alkaline radioactive waste after ruthenium 106 and antimony 125 removal according to example 4.

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EP22153522.2A 2022-01-14 2022-01-26 Procédé d'élimination de radionucléides de déchets radioactifs aqueux Pending EP4213162A1 (fr)

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Citations (5)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
US4116863A (en) * 1976-03-31 1978-09-26 Commissariat A L'energie Atomique Method of decontamination of radioactive effluents
EP2224354A1 (fr) 2009-02-27 2010-09-01 Research In Motion Limited Système de communications fournissant un classement d'efficacité de notification pour affichage de notification et procédés apparentés
CN105032341B (zh) * 2015-08-28 2018-09-28 中国能源建设集团广东省电力设计研究院有限公司 用于处理含铯、锶、钴废水的无机材料及其制备方法
EP3396677A1 (fr) 2015-12-24 2018-10-31 Ebara Corporation Adsorbant pour antimoine radioactif, iode radioactif et ruthénium radioactif, et procédé de traitement de déchets radioactifs liquides utilisant ledit adsorbant
WO2019134437A1 (fr) * 2018-01-04 2019-07-11 清华大学 Adsorbant particulaire de sb2o5, son procédé de préparation et son utilisation pour élimination de 90sr et de 100mag radioactifs

Patent Citations (5)

* Cited by examiner, † Cited by third party
Publication number Priority date Publication date Assignee Title
US4116863A (en) * 1976-03-31 1978-09-26 Commissariat A L'energie Atomique Method of decontamination of radioactive effluents
EP2224354A1 (fr) 2009-02-27 2010-09-01 Research In Motion Limited Système de communications fournissant un classement d'efficacité de notification pour affichage de notification et procédés apparentés
CN105032341B (zh) * 2015-08-28 2018-09-28 中国能源建设集团广东省电力设计研究院有限公司 用于处理含铯、锶、钴废水的无机材料及其制备方法
EP3396677A1 (fr) 2015-12-24 2018-10-31 Ebara Corporation Adsorbant pour antimoine radioactif, iode radioactif et ruthénium radioactif, et procédé de traitement de déchets radioactifs liquides utilisant ledit adsorbant
WO2019134437A1 (fr) * 2018-01-04 2019-07-11 清华大学 Adsorbant particulaire de sb2o5, son procédé de préparation et son utilisation pour élimination de 90sr et de 100mag radioactifs

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